Chemometric Optimization of Solid-Phase Extraction Followed by Liquid Chromatography-Tandem Mass Spectrometry and Probabilistic Risk Assessment of Ultraviolet Filters in an Urban Recreational Lake

1 Introduction

Ultraviolet filters (UVF) are used to protect the human skin from harmful UV radiation and are added to various skin treatment products (Kunze et al., 2021; Kwon and Choi, 2021). However, some UVFs, especially if applied in large quantities, can cause side effects, such as various allergies, dermatitis, and adverse effects on hormonal receptors, nervous system, and reproductive functions (Huang et al., 2021).

Concentrations of individual UVFs in sunscreen preparations are at the level of several percent, and the European Commission (EC No 1223, 2009) has set limit/reference values for individual organic UVFs in the range of 2%–10% (except for drometrizole trisiloxane 15%). UVFs are used daily, and their use is exceptionally high during the summer months (Fagervold et al., 2019), which leads to the release of vast amounts of these substances into the environment (Ma et al., 2016).

Unfortunately, UVFs have been proved to pose a high risk for many aquatic organisms (Carve et al., 2021). Different UVFs affect the environment differently (Labille et al., 2020). Some UVFs tend to accumulate in living cells, affecting reproduction, and increasing mortality in benthic organisms, small fish, and sizeable newborn fish (Carve et al., 2021). This suggests that the presence of UVFs in the water should be considered with great concern.

A significant proportion of UVFs enters the environment through sewage effluents (Wang et al., 2021), which may further contaminate the surface water and groundwater (Li et al., 2020a). In addition, one of the ways of polluting the environment water with UVFs is rinsing the skin during swimming (Teo et al., 2015). Therefore, the presence of UVF needs to be investigated in water at the wastewater treatment plants and in the vicinity of beaches.

Numerous studies have been recently conducted on the occurrence and fate of UVFs in coastal aquatic systems, such as seawater and wastewater (Cadena-Aizaga et al., 2022), corals (Tashiro and Kameda, 2013; Mitchelmore et al., 2021), surface water (Kameda et al., 2011; Tsui et al., 2014), marine water and sediment (Sánchez Rodríguez et al., 2015; Allinson et al., 2018; Mitchelmore et al., 2019), lake sediments (Kaiser et al., 2012), beach sediments (Astel et al., 2020), river sediment (Huang et al., 2016), and fish (Balmer et al., 2005).

Sava Lake in Belgrade (Serbia) is a typical urban lake that is used for recreation such as swimming, sailing, fishing, and diving. In the summer months, there are several thousand people at the lake daily, and it is expected that a large amount of UVFs will be released into the lake water. However, the recreational activities are not evenly distributed along the lake, i.e., there are parts of the lake where there is a big crowd with people sunbathing and swimming and parts of the lake without such activities. Consequently, the different spatial distribution of potential water contaminants is expected.

Risk assessment studies have shown an increased ecological risk due to UVFs in recreational locations and that it depends on the intensity of application of sunscreen products (Teo et al., 2015). Keeping in mind that the concentrations of different UVFs in waters are different and each UVF has a different distribution, the probabilistic approach to risk assessment in swimming water has recently become irreplaceable (Astuti et al., 2022; Dehghani et al., 2022). Compared to the deterministic one, this approach gives a complete picture of the risk estimate, considering that individual UVFs concentrations differ temporarily and spatially (Tsui et al., 2015). In addition to the distribution of UVF concentrations, the distribution of the exposure parameters influencing the risks should not be neglected.

Several analytical methods can be used to quantify the UVFs traces in water. When UVF concentrations are very low, the most optimal technique for sample preparation is solid-phase extraction (SPE) (Allinson et al., 2018; Cadena-Aizaga et al., 2020). This technique enables high degrees of preconcentration, which is why it is the most commonly used technique for analyzing trace level organics in water. In order to get the best analytical performance, the SPE process needs to be optimized (Silva et al., 2013; Chávez-Moreno et al., 2018). As for the instrumental measurement itself, two techniques are predominantly used to measure UVFs. One is gas chromatography with tandem mass spectrometry (GC-MS/MS) (da Silva et al., 2015; Huang et al., 2016; Ramos et al., 2019), which has a huge potential for identification and selectivity in separation. Another technique is liquid chromatography with tandem mass spectrometry (LC-MS/MS) (Li et al., 2020b; Chiriac et al., 2020; Cadena-Aizaga et al., 2022), which is characterized by exceptional sensitivity and is very suitable for the analysis of low-volatile and degradable UVFs.

The main objectives of this work were to optimize the SPE sample preparation prior to LC-MS/MS, investigate the occurrence and spatial distribution of different UVFs in recreational water of an urban city lake, and assess potential environmental risk using a probabilistic approach.

2 Material and Methods

2.1 Study Area and Sampling

The Sava Lake (Figure 1), better known as Ada Ciganlija, is a tributary of the Sava River. The lake was formed about 50 years ago. The length of the lake is about 4.4 km, the average width is 250 m, and the average depth is 4.5 m (Trbojević et al., 2021). The lake volume is about 4 million m³, and the area is approximately 1.0 km². On the left side, there is a small fenced pool connected to the Sava River, from which water is pumped into the Sava Lake, while on the right side, water is discharged from the lake into the Čukarica stream. This artificially ensures water flows through the lake.

FIGURE 1

FIGURE 1. Sampling location - Sava Lake (Serbia).

Sampling was performed in a one-time sampling campaign conducted in August 2021, at the peak of the recreational season. The population of swimmers/bathers on Sava Lake at the time of sampling was about a thousand people. A total of 28 grab samples were taken along the coast and in the middle of Sava Lake. The samples were taken 10 cm below the water surface, stored at 4 °C, and analyzed within 24 h. All water samples were collected in amber glass bottles (volume 0.5 L). Prior to the LC-MS/MS measurement, all samples were subjected to SPE on Oasis^® HLB 6 ml Vac Cartridges with 100 mg sorbent per cartridge (Waters Corp., Milford, MA, United States).

2.2 Sample Preparation

A two-step statistical approach was employed to optimize several variables that affect the SPE sample preparation of UVFs. The variables, such as the type of eluent, percentage of methanol in the rinsing solution (%MeOH), initial pH value, the sample volume (V_s), the rinsing solution volume (V_r), and eluent volume (V_e), were screened by applying Plackett–Burman design (PBD) and were optimized further by central composite design (CCD). The variable and their coded values for PBD are listed in Table 1. PBD experiments, consisting of 15 runs, have been performed according to Supplementary Tables S1, S2, while the subsequent CCD experimental runs are listed in Supplementary Table S3.

TABLE 1

TABLE 1. Plackett-Burman design values for SPE variables.

The effect of pH on the UVFs extraction from sample solution was studied within the range of 2–8, using 0.1 M HCl and 0.1 M NaOH for pH adjustment. Spiked samples were made by dissolving standard mixture solutions of 1.0 μg/ml each UVF in water. After adjusting the initial pH values of the samples, the conditioning of the SPE cartridge was started. A 5 ml volume of the eluent was applied to the cartridges, followed by 5 ml of deionized water whose pH was adjusted to the same value as the pH of the sample to be applied. The sample application was made at approximately 1.0 ml/min flow rate. After applying the sample, the cartridges were washed with a rinsing solution and dried for 10 min. The elution was performed with the selected type of the eluent and its optimized volume. The eluted extracts were evaporated under a stream of nitrogen and reconstituted with 0.5 ml of methanol. All samples were filtered with a 0.22 μm PTFE syringe filter.

2.3 Liquid Chromatography-Tandem Mass Spectrometry Measurement

A Thermo Fisher Scientific (Waltham, United States) LC-MS/MS system comprised of a Dionex Ultimate 3000 liquid chromatograph fitted with an Accucore™ aQ C-18 column (10 cm length, 2.1 mm I.D., particle size 2.6 µm) and LTQ XL linear ion trap mass spectrometer operating in the electrospray ionization (ESI) mode. Mass spectra of analytes were processed by an Xcalibur Ver. 3.0 software. A 10 µL volume of the SPE prepared extract was injected into the LC-MS/MS system. LC mobile phase composition and MS/MS operating parameters are given in Supplementary Tables S4, S5.

2.4 Data Analysis

First, the experimental results were processed by descriptive statistics, Pearson correlation, and the Ryan-Joiner normality test. Then, the log-transformed concentration data were subjected to hierarchical cluster analysis (HCA) using Ward linkage and Euclidean distance. Finally, geostatistical distribution analysis was based on the ordinary kriging method, and results were mapped in the polygon representing Sava Lake.

The ecological risk associated with UVFs in the Sava Lake was assessed based on the risk quotient (RQ), which is the ratio between a measured concentration (C) and a predicted no-effect concentration (PNEC), as described in Eq. 1:

${\displaystyle \sum RQ}={\displaystyle \sum _{i=1}^n\left(C_i/PNE{C}_i\right)}(1)$

Human exposure to UVFs through ingestion and dermal pathways has been evaluated by following the US EPA SWIMODEL exposure assessment model (Li et al., 2020b; Dehghani et al., 2022). Accordingly, the calculation formulas are given in Eqs 2, 3, while the exposure parameters and their values used for risk assessment are listed in Table 2 and Supplementary Tables S6, S7.

$D_{ing}=\left(C_i\cdot IR\cdot ST\cdot SF\cdot BI\right)/\left(AT\cdot BW\right)(2)$

$D_{derm}=\left(DA\cdot SA\cdot SF\right)/\left(AT\cdot BW\right)(3)$

TABLE 2

TABLE 2. Parameters and values used for risk assessment.

Monte Carlo simulation and sensitivity analysis have been made with the following run preferences: the number of trials is 1000, the confidence level is 95%, and the initial seed value of 999.

3 Results and Discussion

3.1 Optimization of SPE of Ultraviolet Filters From Water

3.1.1 Plackett–Burman Design Screening

Since all UVFs are simultaneously subjected to the SPE process, additional efforts should be made to obtain an optimal response that would include all individual responses. Thus, considering that we have 11 UVFs, an aggregate response that includes the individual responses for all analytes simultaneously is used here.

The most commonly used cumulative response in analytical measurements is the desirability function (D) proposed by Derringer and Suich (1980), which represents the geometric mean estimated as a product of the individual desirabilities (d_i) weighted by their individual coefficients (r_i) (Eq. 4). In this case, no difference in weights for individual responses was assumed, so the D values were calculated taking into account all UVFs equally. Therefore, the values for d_i have been maximized and ranged from 0 to 1, while the r_i values were fixed (r_i = 1).

$D={\left({\displaystyle \prod _{i=1}^n{d}_i^{ri}}\right)}^{1/{\displaystyle \sum ri}}(4)$

The results of the screening design are given in the form of a Pareto plot in Figure 2. It shows that the parameter of the most significant influence is the type of SPE eluting solvent. Besides, a considerable influence is also noticed for %MeOH and pH, while other parameters have much less impact on the SPE process. The main effects plot for the tested analytes (Supplementary Figure S1) revealed that in addition to the type of solvent, recoveries are positively affected by increasing the parameters V_e and V_s. Conversely, the increase in the values of the parameters %MeOH, pH, and V_r affect the response negatively.

FIGURE 2

FIGURE 2. Pareto plot of PBD screening SPE variables.

In the second step, ethyl acetate (EtOAc) was selected as an eluent, and the percentage of methanol (%MeOH) in the rinsing solvent and the sample pH value were selected as variables for the CCD optimization.

3.1.2 Central Composite Design Optimization

The initial pH of the sample and %MeOH have been optimized according to CCD in the experimental domain for pH = 2–8 and %MeOH = 2%–8%. Figure 3 shows the response surface plot for optimization of pH and %MeOH. The response was fitted to a second-order polynomial model represented by the following regression equation:

$D=-1.239+0.404\cdot pH+0.362\cdot \%MeOH-0.007\cdot pH\cdot \%MeOH-0.036\cdot p{H}^2-0.034\cdot \%MeO{H}^2(5)$

FIGURE 3

FIGURE 3. Response surface plot of CCD optimization of UVFs.

Final SPE conditions were obtained by optimizing the D value (Figure 3). As a result, a maximum D value of 0.67 was obtained for %MeOH of 4.8% and pH = 5.1. Finally, the global optimum for SPE of all UVFs was selected for the following values of variables: the extraction volume of 150 ml of aqueous sample, pH of the sample set at 5.1, and 15 ml aqueous solution with 4.8%MeOH to rinse the cartridge, and 15 ml EtOAc for elution. These conditions were used to prepare water samples from Sava Lake for the analysis of UVFs by the LC-MS/MS method.

3.2 Validation of SPE-LC-MS/MS Method

The optimized SPE sample preparation was accompanied by LC-MS/MS measurement. The LC-MS/MS method was previously optimized, which included optimizing the HPLC mobile phase (Vasiljević et al., 2004), tuning the MS instrument, finding optimal m/z and values, and CID value optimization (Grujić et al., 2009). The optimal LC-MS/MS parameters are given in Supplementary Tables S4, S5. Typical LC-MS/MS chromatograms for eleven UVFs detected in Sava Lake water are shown in Figure 4. Supplementary Figures S2–S31 present the LC-MS/MS chromatograms for all samples, blank and a standard mixture.

FIGURE 4

FIGURE 4. LC-MS/MS chromatograms of UVFs in a real water sample (no. 20) from Sava Lake.

In order to assess the analytical performances of the method, the method detection limits (MDL), average recovery (R), and relative standard deviation (RSD) were determined. Clean surface water, in which the analyzed UVFs were not detected, was used to make spiked samples and construct matrix-matched calibration lines at nine concentration levels for the UVFs mixture. The calibration range was 0.1–300 ng/L. For each UVF, the linear correlation coefficient was greater than 0.995. The obtained MDL, R, and RSD values are listed in Supplementary Table S8. MDLs, estimated as three times the signal-to-noise ratio, range from 0.01 to 4.4 ng/L. Recovery studies were performed at 1.0, 10, and 100 ng/L concentration levels. Average recoveries for 11 analytes range from 44% to 99%. Six replicates were used to investigate repeatability at the mentioned concentration levels, and RSDs values within ±19% were obtained.

3.3 Occurrence of Ultraviolet Filters in Recreational Lake Water

Descriptive statistics, along with the distribution parameters, are presented in Table 3. The concentration profile of most of the tested UVFs in the studied Sava Lake shows a log-normal distribution skewed to the right, which is shown by positive values for skewness. All skewness values are greater than 1.0, except for BP-1, BP-3, and 4-HB. These three UVFs have negative kurtosis, indicating platykurtic distributions, i.e., flatter tails. Mean values of UVFs substances in the investigated water were different in different parts of the lake. The obtained concentrations range from 0.09 ng/L for IAMC to 584 ng/L for EHMC. The highest average concentration was detected for EHMC at 113 ng/L, and the least present UVFs detected were IAMC and OD-PABA, with average concentrations of 0.3 ng/L and 0.4 ng/L, respectively. These two UVFs were detected only in parts of the lake where human recreational activity (swimming/bathing) is intense, while the other nine UVFs were detected in all samples. Total mean concentrations of UVFs decrease in the following order: EHMC > 4-MBC > BP-3 > OC > AVO > 4-HB > HMS > BP-4 > BP-1 > OD-PABA > IAMC.

TABLE 3

TABLE 3. Descriptive statistics of UVFs in Sava Lake (ng/L).

The content of these UVFs in Sava Lake water varies significantly, so it is somewhat inconvenient to compare it with other recreational waters. However, one may conclude that the level of concentrations obtained is in the range of concentrations in other cited studies, including coastal marine water: 0.07–172 μg/L (Cadena-Aizaga et al., 2022), n.d.–3730 ng/L, n.d.–1298 ng/L, n.d.–341 ng/L (Kwon and Choi, 2021), swimming pool water: up to 1500 μg/L (Mokh et al., 2021), n.d.–289 ng/L (Li et al., 2020b), lake water: <2–35 ng/L (Balmer et al., 2005), drinking and river water: 44–105 ng/L (da Silva et al., 2015), and municipal wastewater: 0.1–19 μg/L (Balmer et al., 2005), n.d.–400 ng/L (Wang et al., 2021), 621–951 ng/L (Wu et al., 2018).

Pearson correlation matrix (Supplementary Table S9) reveals a strong association between UVFs. Only OD-PABA concentrations are not related to other UVFs. The highest correlation coefficient of 0.969 was found for the pair EHMC and AVO, while the smallest one was estimated for the pair BP-1 and OD-PABA (0.102). In general, it can be concluded that there is a large intercorrelation between UVFs. Figure 5 shows a dendrogram obtained by hierarchical cluster analysis (HCA). The relationship between the groups of tested samples and UVFs is obvious. Four clusters (I, II, III, and IV) were identified. This grouping can be attributed to the different spatial distribution of sampling points and the difference in the amount of UVFs in sunscreen products and how they are applied. Namely, sunscreen products are usually composed of a combination of UVFs to ensure the broadest protection.

FIGURE 5

FIGURE 5. Dendrogram of water samples from Sava Lake.

3.4 Environmental Risk Assessment

3.4.1 Deterministic Approach

RQs for individual UVFs were obtained by dividing C_i obtained in this study by PNECs values (Supplementary Table S10), which are collected after the literature survey (Lukić et al., 2021). The risk classification was based on risk ranking criteria in which RQ < 0.01; 0.01 < RQ < 0.1; 0.1 < RQ < 1; and RQ > 1, are “Unlikely to pose risk”; “Low risk”; “Medium risk” and “High risk”, respectively (Ma et al., 2016).

Contributions of individual UVFs to total RQ are presented in Figure 6. It is noticeable that the greatest contribution to RQ is made by the presence of EHMC, followed by 4-MBC and BP-1. The share of other UVFs in total RQ can be almost neglected. The estimated minimum, average and maximum RQs values are 0.4, 0.35 and 1.7, respectively. There are two groups of samples in which the RQ values exceed 1. The first group comprises samples that highly exceed one and are marked 13–15, while the second group includes samples numbered 12, 27, and 28, slightly above 1. In conclusion, both sample groups represent locations with a high ecological risk.

FIGURE 6

FIGURE 6. Contribution of individual UVFs to total RQ.

The geostatistical distribution of risk in Sava Lake was made based on calculated RQs from the measured values, which were used to perform ordinary kriging interpolation on the entire lake area (Radomirović et al., 2020). Figure 7 shows that in several places close to the lake beach, the RQs are elevated in comparison to the middle of the lake. Several hotspots have been identified (A, B, C, D), which correlate with the intensity of human activities at the site.

FIGURE 7

FIGURE 7. Geostatistical distribution of ΣRQ in Sava Lake.

In area A, samples 12, 13, 14, and 15 are located, while samples 27 and 28 are in area B. These samples show RQ ˃ 1 (Figure 6) and are classified in clusters III and IV in the dendrogram (Figure 5). Samples 19 and 20 are in area D, and sample 22 represents sampling point C. This distribution reflects the intensity of human activity at the lake. Most people and swimmers/bathers are located on the beach and in the water in area A, then an area at point B. At locations C and D, there are beaches with significantly fewer people. In the middle of the lake, as well as at the left and right edges, water contamination with UVFs is significantly lower.

3.4.2 Monte Carlo Simulation and Sensitivity Analysis

Since UVFs concentrations are not uniformly distributed across the lake, a probabilistic approach to human exposure is expected to provide a more realistic assessment than a point estimate (Astuti et al., 2022; Dehghani et al., 2022). Given that the exposure parameters also have their distributions, individual risks and cumulative risk will also follow some distributions. Namely, the exposure parameters AT and BI are fixed points, SF and ST have triangle distribution, while BW and SA follow a log-normal distribution. PNEC, Log Kow, and MW are analyte-specific fixed-values (Table 2, Supplementary Tables S6, S7). Concentrations of individual UVFs have been fitted to estimate the best distribution. All UVFs concentrations follow a log-normal distribution, except BP-4, which is best fitted with the Webuill curve.

Monte Carlo simulation of human exposure was applied to UVFs in Sava Lake. According to the SWIMMER model, humans may be exposed to UVFs through inhalation, digestion, and dermal pathway. While inhalation is less likely to be a significant route due to the low volatility of UVFs (Lu et al., 2017), the other two are expected to be the important exposure routes of UVFs to humans. The accidental ingestion and dermal absorption of UVFs were calculated from Eqs 2, 3. The exposure parameters listed in Table 2 were used to estimate the human dose for adults and children (age 11–14 years). The Monte Carlo calculation results are presented in Supplementary Table S11.

Human exposure through the dermal pathway poses a higher risk compared to ingestion for most UVFs, except for BP-1, BP-3, BP-4 and 4-HB. Figure 8 shows the human exposure distribution for adults and children and the corresponding sensitivity risk analysis. The histograms for the total exposure dose show the simulated ΣD_a and ΣD_c in 90% (the 90 of the estimated percentile) for the adult and children groups of 47.5 and 77.5 ng/kg∙day, respectively. This indicates that children are much more at risk due to UVFs exposure than adults because of their lower body-weight/skin surface ratio. Anyway, the lack of reference dose (R_fD) values prevents the explicit expression of the health risk index. Instead, the UVFs exposure can be compared to similar substances, i.e., parabens for which there is R_fD of 10 mg/kg∙BW/day (Li et al., 2021) proposed by the Joint Expert Committee on Food Additives (JECFA) of Food and Agriculture Organization of the United Nations (FAO) and World Organization (WHO). Based on this comparison, it can be concluded that there is a negligible risk to human health for the estimated UVFs doses (ng/kg∙day) (Li et al., 2020B). Thus, the concentrations of these compounds in Sava Lake water can be considered acceptable, except at a few hotspot locations. Anyhow, there are concerns that UVFs will affect human health in the long term either through their influence or from harmful organic substances that may arise as products of their degradation.

FIGURE 8

FIGURE 8. Probability and sensitivity analysis of different groups exposed to UVFs: (A) adults; (B) children.

4 Conclusion

SPE may be efficiently step-wise optimized using screening and response surface designs. It is a reliable sample preparation technique, which, coupled with LC-MS/MS, represents a suitable analytical tool for UVFs in surface water. Among 11 popular UVFs, EHMC, 4-MBC, and BP-3 were most abundant in the studied recreational lake. It was shown that recreational activities greatly influenced the occurrence of UVFs, their spatial distribution, and potential environmental risk. UVFs are significantly present near the coast, i.e., close to the beach. Nevertheless, the RQ values exceeded one at several locations in the lake. The incidental ingestion is a minor route to human exposure to most UVFs. Monte Carlo simulation of risk estimated 63% higher percentiles for total human exposure of children compared to adults. In addition, the sensitivity identified the most influential variables as the content of EHMC, HMS, and 4-MBC, along with two exposure parameters, human body weight and skin surface area. In general, except for the high ecological risk in some parts of the lake, UVFs in studied recreational lake water posed no concern to human health in the short term.

Data Availability Statement

The original contributions presented in the study are included in the article/Supplementary Material, further inquiries can be directed to the corresponding author.

Author Contributions

JL: methodology, investigation, and writing–original draft. JR: resources and validation. ML: formal analysis and visualization. TĐ: supervision, project administration, and funding acquisition. AO: conceptualization, software, writing–review and editing.

Funding

This research was supported by the Ministry of Education, Science and Technological Development of the Republic of Serbia (Grants 451-03-68/2022-14/200287 and 451-03-68/2022-14/200135).

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Publisher’s Note

All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors, and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.

Supplementary Material

The Supplementary Material for this article can be found online at: https://www.frontiersin.org/articles/10.3389/fenvs.2022.916916/full#supplementary-material

References

Allinson, M., Kameda, Y., Kimura, K., and Allinson, G. (2018). Occurrence and Assessment of the Risk of Ultraviolet Filters and Light Stabilizers in Victorian Estuaries. Environ. Sci. Pollut. Res. 25, 12022–12033. doi:10.1007/s11356-018-1386-7

CrossRef Full Text | Google Scholar

Astel, A., Stec, M., and Rykowska, I. (2020). Occurrence and Distribution of UV Filters in Beach Sediments of the Southern Baltic Sea Coast. Water 12, 3024. doi:10.3390/w12113024

CrossRef Full Text | Google Scholar

Astuti, R. D. P., Mallongi, A., Choi, K., Amiruddin, R., Hatta, M., Tantrakarnapa, K., et al. (2022). Health Risks from Multiroute Exposure of Potentially Toxic Elements in a Coastal Community: A Probabilistic Risk Approach in Pangkep Regency, Indonesia. Geomatics, Nat. Hazards Risk 13, 705–735. doi:10.1080/19475705.2022.2041110

CrossRef Full Text | Google Scholar

Balmer, M. E., Buser, H.-R., Müller, M. D., and Poiger, T. (2005). Occurrence of Some Organic UV Filters in Wastewater, in Surface Waters, and in Fish from Swiss Lakes. Environ. Sci. Technol. 39, 953–962. doi:10.1021/es040055r

PubMed Abstract | CrossRef Full Text | Google Scholar

Cadena-Aizaga, M. I., Montesdeoca-Esponda, S., Torres-Padrón, M. E., Sosa-Ferrera, Z., and Santana-Rodríguez, J. J. (2020). Organic UV Filters in Marine Environments: An Update of Analytical Methodologies, Occurrence and Distribution. Trends Environ. Anal. Chem. 25, e00079. doi:10.1016/j.teac.2019.e00079

CrossRef Full Text | Google Scholar

Cadena-Aizaga, M. I., Montesdeoca-Esponda, S., Sosa-Ferrera, Z., and Santana-Rodríguez, J. J. (2022). Occurrence and Environmental Hazard of Organic UV Filters in Seawater and Wastewater from Gran Canaria Island (Canary Islands, Spain). Environ. Pollut. 300, 118843. doi:10.1016/j.envpol.2022.118843

PubMed Abstract | CrossRef Full Text | Google Scholar

Carve, M., Nugegoda, D., Allinson, G., and Shimeta, J. (2021). A Systematic Review and Ecological Risk Assessment for Organic Ultraviolet Filters in Aquatic Environments. Environ. Pollut. 268, 115894. doi:10.1016/j.envpol.2020.115894

PubMed Abstract | CrossRef Full Text | Google Scholar

Chávez-Moreno, C. A., Hinojosa-Reyes, L., Ruiz-Ruiz, E. J., Hernández-Ramírez, A., and Guzmán-Mar, J. L. (2018). Optimization of Solid-phase Extraction of Parabens and Benzophenones in Water Samples Using a Combination of Plakett-Burman and Box-Behnken Designs. J. Sep. Sci. 41, 4488–4497. doi:10.1002/jssc.201800796

PubMed Abstract | CrossRef Full Text | Google Scholar

Chiriac, F. L., Paun, I., Pirvu, F., Pascu, L. F., Niculescu, M., and Galaon, T. (2020). Liquid Chromatography Tandem Mass Spectrometry Method for Ultra-trace Analysis of Organic UV Filters in Environmental Water Samples. Rev. Chim. 71, 92–99. doi:10.37358/RC.20.1.7818

CrossRef Full Text | Google Scholar

da Silva, C. P., Emídio, E. S., and de Marchi, M. R. R. (2015). The Occurrence of UV Filters in Natural and Drinking Water in São Paulo State (Brazil). Environ. Sci. Pollut. Res. 22, 19706. doi:10.1007/s11356-015-5174-3

CrossRef Full Text | Google Scholar

Dehghani, M., Shahsavani, S., Mohammadpour, A., Jafarian, A., Arjmand, S., Rasekhi, M. A., et al. (2022). Determination of Chloroform Concentration and Human Exposure Assessment in the Swimming Pool. Environ. Res. 203, 111883. doi:10.1016/j.envres.2021.111883

PubMed Abstract | CrossRef Full Text | Google Scholar

Derringer, G., and Suich, R. (1980). Simultaneous Optimization of Several Response Variables. J. Qual. Technol. 12, 214–219. doi:10.1080/00224065.1980.11980968

CrossRef Full Text | Google Scholar

EC No 1223, (2009). Regulation (EC) No 1223/2009 of the European Parliament and of the Council of 30 November 2009 on Cosmetic Products. Official Journal of the European Union L. 342, 59.

Google Scholar

Fagervold, S. K., Rodrigues, A. S., Rohée, C., Roe, R., Bourrain, M., Stien, D., et al. (2019). Occurrence and Environmental Distribution of 5 UV Filters during the Summer Season in Different Water Bodies. Water. Air. Soil Pollut. 230, 172. doi:10.1007/s11270-019-4217-7

CrossRef Full Text | Google Scholar

Grujić, S., Vasiljević, T., and Laušević, M. (2009). Determination of Multiple Pharmaceutical Classes in Surface and Ground Waters by Liquid Chromatography-Ion Trap-Tandem Mass Spectrometry. J. Chromatogr. A 1216, 4989–5000. doi:10.1016/j.chroma.2009.04.059

PubMed Abstract | CrossRef Full Text | Google Scholar

Huang, W., Xie, Z., Yan, W., Mi, W., and Xu, W. (2016). Occurrence and Distribution of Synthetic Musks and Organic UV Filters from Riverine and Coastal Sediments in the Pearl River Estuary of China. Mar. Pollut. Bull. 111, 153–159. doi:10.1016/j.marpolbul.2016.07.018

PubMed Abstract | CrossRef Full Text | Google Scholar

Huang, Y., Law, J. C.-F., Lam, T.-K., and Leung, K. S.-Y. (2021). Risks of Organic UV Filters: a Review of Environmental and Human Health Concern Studies. Sci. Total Environ. 755, 142486. doi:10.1016/j.scitotenv.2020.142486

PubMed Abstract | CrossRef Full Text | Google Scholar

Kaiser, D., Wappelhorst, O., Oetken, M., and Oehlmann, J. (2012). Occurrence of Widely Used Organic UV Filters in Lake and River Sediments. Environ. Chem. 9, 139. doi:10.1071/EN11076

CrossRef Full Text | Google Scholar

Kameda, Y., Kimura, K., and Miyazaki, M. (2011). Occurrence and Profiles of Organic Sun-Blocking Agents in Surface Waters and Sediments in Japanese Rivers and Lakes. Environ. Pollut. 159, 1570–1576. doi:10.1016/j.envpol.2011.02.055

PubMed Abstract | CrossRef Full Text | Google Scholar

Kunze, G., Schlifke, A., Jackson, E., Hefner, N., Berg, K., and Vollhardt, J. (2021). A Novel, Benchmark-Centered, Eco-Impact Rating System for Sunscreens and Sunscreen Formulation Design. Front. Environ. Sci. 9, 727404. doi:10.3389/fenvs.2021.727404

CrossRef Full Text | Google Scholar

Kwon, B., and Choi, K. (2021). Occurrence of Major Organic UV Filters in Aquatic Environments and Their Endocrine Disruption Potentials: A Mini‐review. Integr. Environ. Assess Manag. 17, 940–950. doi:10.1002/ieam.4449

PubMed Abstract | CrossRef Full Text | Google Scholar

Labille, J., Catalano, R., Slomberg, D., Motellier, S., Pinsino, A., Hennebert, P., et al. (2020). Assessing Sunscreen Lifecycle to Minimize Environmental Risk Posed by Nanoparticulate UV-Filters - A Review for Safer-By-Design Products. Front. Environ. Sci. 8, 101. doi:10.3389/fenvs.2020.00101

CrossRef Full Text | Google Scholar

Li, X., Tian, T., Shang, X., Zhang, R., Xie, H., Wang, X., et al. (2020a). Occurrence and Health Risks of Organic Micro-pollutants and Metals in Groundwater of Chinese Rural Areas. Environ. Health Perspect. 128, 107010. doi:10.1289/EHP6483

PubMed Abstract | CrossRef Full Text | Google Scholar

Li, Y., Chen, L., Li, H., Peng, F., Zhou, X., and Yang, Z. (2020b). Occurrence, Distribution, and Health Risk Assessment of 20 Personal Care Products in Indoor and Outdoor Swimming Pools. Chemosphere 254, 126872. doi:10.1016/j.chemosphere.2020.126872

PubMed Abstract | CrossRef Full Text | Google Scholar

Li, C., Zhao, Y., Liu, S., Yang, D., Ma, H., Zhu, Z., et al. (2021). Exposure of Chinese Adult Females to Parabens from Personal Care Products: Estimation of Intake via Dermal Contact and Health Risks. Environ. Pollut. 272, 116043. doi:10.1016/j.envpol.2020.116043

PubMed Abstract | CrossRef Full Text | Google Scholar

Lu, J., Mao, H., Li, H., Wang, Q., and Yang, Z. (2017). Occurrence of and Human Exposure to Parabens, Benzophenones, Benzotriazoles, Triclosan and Triclocarban in Outdoor Swimming Pool Water in Changsha, China. Sci. Total Environ. 605-606, 1064–1069. doi:10.1016/j.scitotenv.2017.06.135

PubMed Abstract | CrossRef Full Text | Google Scholar

Lukić, J., Rvović, S., Đurkić, T., and Onjia, A. (2021). Procena Ekološkog Rizika Usled Prisustva Organskih UV Filtera U Vodi I Sedimentima. Ecologica 28, 325–330. doi:10.18485/ecologica.2021.28.102.26

CrossRef Full Text | Google Scholar

Ma, B., Lu, G., Liu, F., Nie, Y., Zhang, Z., and Li, Y. (2016). Organic UV Filters in the Surface Water of Nanjing, China: Occurrence, Distribution and Ecological Risk Assessment. Bull. Environ. Contam. Toxicol. 96, 530–535. doi:10.1007/s00128-015-1725-z

PubMed Abstract | CrossRef Full Text | Google Scholar

Mitchelmore, C. L., He, K., Gonsior, M., Hain, E., Heyes, A., Clark, C., et al. (2019). Occurrence and Distribution of UV-Filters and Other Anthropogenic Contaminants in Coastal Surface Water, Sediment, and Coral Tissue from Hawaii. Sci. Total Environ. 670, 398–410. doi:10.1016/j.scitotenv.2019.03.034

PubMed Abstract | CrossRef Full Text | Google Scholar

Mitchelmore, C. L., Burns, E. E., Conway, A., Heyes, A., and Davies, I. A. (2021). A Critical Review of Organic Ultraviolet Filter Exposure, Hazard, and Risk to Corals. Environ. Toxicol. Chem. 40, 967–988. doi:10.1002/etc.4948

PubMed Abstract | CrossRef Full Text | Google Scholar

Mokh, S., Nassar, R., Berry, A., Doumiati, S., Taha, M., Ezzeddine, R., et al. (2021). Chromatographic Methods for the Determination of a Broad Spectrum of UV Filters in Swimming Pool Water. Environ. Sci. Pollut. Res. 29, 18605–18616. doi:10.21203/rs.3.rs-284258/v1

CrossRef Full Text | Google Scholar

Radomirović, M., Ćirović, Ž., Maksin, D., Bakić, T., Lukić, J., Stanković, S., et al. (2020). Ecological Risk Assessment of Heavy Metals in the Soil at a Former Painting Industry Facility. Front. Environ. Sci. 8, 560415. doi:10.3389/fenvs.2020.560415

CrossRef Full Text | Google Scholar

Ramos, S., Homem, V., and Santos, L. (2019). Simultaneous Determination of Synthetic Musks and UV-Filters in Water Matrices by Dispersive Liquid-Liquid Microextraction Followed by Gas Chromatography Tandem Mass-Spectrometry. J. Chromatogr. A 1590, 47–57. doi:10.1016/j.chroma.2019.01.013

PubMed Abstract | CrossRef Full Text | Google Scholar

Sánchez Rodríguez, A., Rodrigo Sanz, M., and Betancort Rodríguez, J. R. (2015). Occurrence of Eight UV Filters in Beaches of Gran Canaria (Canary Islands). An Approach to Environmental Risk Assessment. Chemosphere 131, 85–90. doi:10.1016/j.chemosphere.2015.02.054

PubMed Abstract | CrossRef Full Text | Google Scholar

Silva, C. P. D., Emídio, E. S., and Marchi, M. R. R. D. (2013). UV Filters in Water Samples: Experimental Design on the SPE Optimization Followed by GC-MS/MS Analysis. J. Braz. Chem. Soc. 24, 1433. doi:10.5935/0103-5053.20130182

CrossRef Full Text | Google Scholar

Tashiro, Y., and Kameda, Y. (2013). Concentration of Organic Sun-Blocking Agents in Seawater of Beaches and Coral Reefs of Okinawa Island, Japan. Mar. Pollut. Bull. 77, 333–340. doi:10.1016/j.marpolbul.2013.09.013

PubMed Abstract | CrossRef Full Text | Google Scholar

Teo, T. L. L., Coleman, H. M., and Khan, S. J. (2015). Chemical Contaminants in Swimming Pools: Occurrence, Implications and Control. Environ. Int. 76, 16–31. doi:10.1016/j.envint.2014.11.012

PubMed Abstract | CrossRef Full Text | Google Scholar

Trbojević, I. S., Popović, S. S., Milovanović, V. V., Predojević, D. D., Subakov Simić, G. V., Jakovljević, O. S., et al. (2021). Substrate Type Selection in Diatom Based Lake Water Quality Assessment. Knowl. Manag. Aquat. Ecosyst. 21, 12. doi:10.1051/kmae/2021022

CrossRef Full Text | Google Scholar

Tsui, M. M. P., Leung, H. W., Wai, T.-C., Yamashita, N., Taniyasu, S., Liu, W., et al. (2014). Occurrence, Distribution and Ecological Risk Assessment of Multiple Classes of UV Filters in Surface Waters from Different Countries. Water Res. 67, 55–65. doi:10.1016/j.watres.2014.09.013

PubMed Abstract | CrossRef Full Text | Google Scholar

Tsui, M. M. P., Leung, H. W., Kwan, B. K. Y., Ng, K.-Y., Yamashita, N., Taniyasu, S., et al. (2015). Occurrence, Distribution and Ecological Risk Assessment of Multiple Classes of UV Filters in Marine Sediments in Hong Kong and Japan. J. Hazard. Mater. 292, 180–187. doi:10.1016/j.jhazmat.2015.03.025

PubMed Abstract | CrossRef Full Text | Google Scholar

Vasiljević, T., Onjia, A., Čokeša, Đ., and Laušević, M. (2004). Optimization of Artificial Neural Network for Retention Modeling in High-Performance Liquid Chromatography. Talanta 64, 785–790. doi:10.1016/j.talanta.2004.03.032

PubMed Abstract | CrossRef Full Text | Google Scholar

Wang, S., Huo, Z., Gu, J., and Xu, G. (2021). Benzophenones and Synthetic Progestin in Wastewater and Sediment from Farms, WWTPs and Receiving Surface Water: Distribution, Sources, and Ecological Risks. RSC Adv. 11, 31766–31775. doi:10.1039/D1RA05333G

PubMed Abstract | CrossRef Full Text | Google Scholar

Wu, M.-h., Li, J., Xu, G., Ma, L.-d., Li, J.-j., Li, J.-s., et al. (2018). Pollution Patterns and Underlying Relationships of Benzophenone-type UV-Filters in Wastewater Treatment Plants and Their Receiving Surface Water. Ecotoxicol. Environ. Saf. 152, 98–103. doi:10.1016/j.ecoenv.2018.01.036

PubMed Abstract | CrossRef Full Text | Google Scholar